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Abstract

Polybrominated diphenyl ethers (PBDEs) were introduced in the late 1970's as additive flame retardants incorporated into textiles, electronics, plastics and furniture. Although 2,2',3,3',4,4',5,5',6,6'-decabromodiphenyl ether (BDE209) is the only congener currently on the market, 2,2`,4,4`-tetrabromodiphenyl ether (BDE47), 2,2`,4,4`,5-pentabromodiphenyl ether (BDE99), and 2,2`,4,4`,5,5`-hexabromodiphenyl ether (BDE153) are the predominant congeners detected in human and wildlife samples. Upon exposure, PBDEs enter the liver where they are biotransformed to potentially toxic metabolites. Although the human liver burden of PBDEs is not clear, the presence of PBDEs in human liver is particularly alarming because it has been demonstrated in rodents that hydroxylated metabolites may play a pivotal role in PBDE-mediated toxicity. The mechanism by which PBDEs enter the liver was not known. However, due to their large molecular weights (MWs ~485 to 1000 Da), they were not likely to enter hepatocytes by simple diffusion. Organic anion transporting polypeptides (OATPs: human; Oatps: rodents) are responsible for hepatic uptake of a variety of amphipathic compounds of MWs larger than 350 Da. Therefore, I tested the hypothesis that OATPs/Oatps expressed in human and mouse hepatocytes are responsible for the uptake of PBDE congeners 47, 99, and 153 by using Chinese hamster ovary (CHO) cell lines expressing OATP1B1, OATP1B3, or OATP2B1 and Human Embryonic Kidney 293 (HEK293) cells transiently expressing Oatp1a1, Oatp1a4, Oatp1b2, or Oatp2b1. Direct uptake studies illustrated that PBDE congeners are substrates of human and mouse hepatic OATPs/Oatps, except for Oatp1a1. Detailed kinetic analysis revealed that OATP1B1, OATP1B3, Oatp1a4, and Oatp1b2 transport BDE47 with the highest affinity followed by BDE99 and BDE153. However, both OATP2B1 and Oatp2b1 transported all three congeners with similar affinities. The importance of hepatic Oatps for the accumulation of BDE47 in liver was confirmed using Oatp1a4- and Oatp1b2-null mice. These results clearly suggest that uptake of PBDEs via these OATPs/Oatps are responsible for liver-specific accumulation of PBDEs. In mouse liver, PBDEs induce drug metabolizing enzymes, namely cytochrome P450s (Cyps). However, the molecular mechanisms underlying this induction was unknown. Cyp2b10 and 3a11 are target genes of the xenobiotic nuclear receptors, the constitutive androstane receptor (CAR) and pregnane X receptor (PXR), both of which are responsible for mediating induction of Cyp2b10 and Cyp3a11, respectively. I hypothesized that PBDE congeners are CAR and/or PXR activators. Using reporter-gene luciferase assays I showed that BDE47, BDE99 and BDE209 activate human and mouse CAR and PXR in a concentration-dependent manner. Furthermore, induction of Cyp2b10 and Cyp3a11 was markedly suppressed in CAR- and PXR-null mice, respectively, indicating that PBDE congeners activate these receptors in vivo. BDE47 and BDE99, the primary congeners detected in humans in the United States, are capable of inducing Cyp2b and Cyp3a enzymes in rodents. However, it is not clear which Cyp isoform, if any, is preferentially induced upon exposure to BDE47 or BDE99. Induction of mouse hepatic Cyp2b10 and 3a11 by PBDEs showed distinct dose-responses, with Cyp2b10 being induced at lower doses and Cyp3a11 at much higher doses, indicating PBDEs are more likely to induce hepatic enzymes at doses that humans are exposured to. Currently, daily exposure of PBDEs is estimated to be 0.003mg/kg for adults. This study shows that effects of PBDEs are seen in animal models at concentrations within ~10-fold of the high end of the human population. Together, the results from the current dissertational study demonstrate that PBDEs are substrates of OATPs/Oatps and activators of CAR and PXR. This study not only provides a molecular basis for understanding PBDE disposition and toxicity in the liver but also cautions PBDE exposure may result in broader impact on liver physiology and toxicology.